Spatial analysis of the benefits and burdens of ecological focus areas for water-related ecosystem services vulnerable to climate change in Europe

There are many concerns regarding the effects of climate change including threats to ecosystem services. Rural land use can influence these services and there is scope for associated policies to steer decisions towards maximising benefits and minimising burdens. In Europe, for example, ecological focus areas (EFAs), introduced in the last reform of the Common Agricultural Policy, can have impacts on ecosystem services which vary with location, including potential trade-offs between benefits and burdens in some regions. This study combines the outputs from two continental-scale projects to provide a new perspective on the potential impact of EFAs for water-related ecosystem services under threat from climate change. An ecosystem service impact indicator framework was applied in conjunction with a climate change vulnerability assessment. This resulted in vulnerability and area weighted performance scores for dilution, filtration, water provision, and flood regulation services for 10 EFAs in 1256 regions. Best, average and worst case scenario maps were created that highlight the relative benefits and burdens of EFAs. Six EFAs have been identified which have not been activated in nine European Member States but which have potential to provide benefits. Eleven Member States have been identified which have regions where 3 EFAs should be avoided due to potential burdens. This analysis facilitates broad spatial targeting on a continental-scale of specific EFAs which may help maintain (and ideally increase) ecosystem service capacity and resilience in vulnerable regions.


Introduction
There are many concerns regarding the potential negative effects of climate change and amongst these are potential threats to ecosystem services such as increases in soil erosion and flooding, decreases in water provision and water quality and a reduction in pollination (Chang and Bonnette 2016;Dunford et al. 2015;Jentsch and Beierkuhnlein 2008;Maron et al. 2017;Lindner et al. 2010;Panagos et al. 2017;Runting et al. 2017;Vanbergen 2013;Wilby et al. 2010). Many of these services are influenced and impacted upon by agricultural land use practices. Consequently, policies that govern these, such as the Common Agricultural Policy (CAP) in Europe, can have benefits and burdens (positive and negative effects and impacts) on ecosystem services within a region, nation, across a whole continent such as Europe, and consequently globally. In the last reform of the CAP in 2013 (EC 2013a, b, c, d), a number of 'greening' measures were introduced, including a requirement for farms with more than 15 ha of arable land to dedicate at least 5% of their arable land to ecological focus areas (EFAs). As the name suggests, EFAs are land use and landscape features that potentially provide ecological benefits. Globally, this could include a broad range of land and features, but in the context of the European CAP it refers to a specific set of 19 land uses and features. The principal objective of these European EFAs is to contribute towards maintaining and enhancing biodiversity (EC 2013c), driven by the historic decline in farmland biodiversity (Chamberlain et al. 2000;Cresswell 2010;Donald et al. 2001;Goulson et al. 2008;Newton 2004;Temple and Terry 2007). However, EFAs may also have benefits for ecosystem services (Tzilivakis et al. 2015b) which have also been subject to declines in recent decades (Harrison et al. 2010;IPBES 2016;MEA 2005;SEP 2015).
The need to address historic and current issues has been at the core of many agrienvironmental policies and measures. However, there is an increasing need to also account for future threats (EEA 2009(EEA , 2011SEP 2016). This includes near future issues, such as emerging pollutants (Brack et al. 2015) or medium-and long-term issues such as climate change. The latter of these is explored within this study, the objective of which was to combine the outputs from two continental-scale projects to provide a new perspective on the potential benefits and burdens of EFAs with respect to addressing climate change threats to waterrelated ecosystem services. An indicator framework to assess the ecosystem service impacts of EFAs (Tzilivakis et al. 2016) is applied in conjunction with an assessment of the vulnerability of ecosystem services to climate change (Tzilivakis et al. 2015a).
The indicator framework was developed to support a software tool, the EFA Calculator (AERU 2017), that aims to identify EFAs for a farm that offer the greatest potential benefits and least burdens. It takes into account numerous farm-specific geographical and management factors to derive performance scores for EFAs, thus steering farms towards selecting those with the highest performance score for their specific circumstances. The assessment of the vulnerability of ecosystem services to climate change was undertaken to support the development of the Optimal Strategies for Climate Change Action in Rural areas (OSCAR) software application (AERU 2013(AERU , 2014. OSCAR aims to assess the climate change mitigation and adaptation benefits and burdens of measures and operations available within the European Rural Development Programme (RDP). The adaptation assessment routines in OSCAR utilise the assessment of the vulnerability of ecosystem services to climate change to provide an assessment of the potential impact of RDP operations.
The overlap in these two projects, with respect to ecosystem services, provides scope to combine them and consequently provide new insights for future land use and management policy. In this study, the outputs of this combining process have been used to identify European regions where particular EFAs may be beneficial with respect to increasing ecosystem service capacity, and consequently increasing resilience and the ability to cope with climate change. This study has been applied in the context of the European continent, but the approaches utilised are sufficiently flexible to be applied to other countries and continents around the world. For example, the indicator framework could be tailored for other land uses and landscape features found outside of Europe and this could then be combined with climate change vulnerability assessments for non-European countries and continents. Additionally, many of the land use and landscape features examined (e.g. afforested areas, agroforestry, buffer strips, ditches, fallow land, ponds, etc.) are utilised elsewhere in the world, so understanding their benefits and burdens in a European context may be valuable when considering their potential impact elsewhere (especially when regional circumstances are similar).

Overview
The EFA Calculator software (AERU 2017; Tzilivakis et al. 2015b) was used to assess the relative benefits and burdens for ecosystem services from different EFAs in each level 3 Nomenclature of Territorial Units for Statistics (NUTS3) region in the European Union (EU). These benefits/burdens were combined with the assessment of the vulnerability of ecosystem services to climate change identified in Tzilivakis et al. (2015a) to facilitate a spatial analysis. This analysis identifies regions where EFAs have the potential to increase the capacity of water-related ecosystem services, taking into account climate change vulnerabilities.
The approach can be broadly split into two steps: 1. Data generation: Creation of the NUTS3 farms (input data) and running this data through the EFA calculator to generate data on potential ecosystem service benefits and burdens for each farm for each EFA. 2. Data analysis: Processing data output from the EFA calculator to account for climate change vulnerabilities, including using geographical information systems (GIS) to visualise the results in a map format. Tzilivakis et al. (2015a) assessed the vulnerability of regions to climate change in relation to nine ecosystem services. This study focuses on the four water-related services of dilution, filtration, flood regulation and water provision. These were selected for two reasons. Firstly, because the spatial attributes that influence the impact of EFAs on these services are likely to vary regionally. Secondly, the other services, such as soil erosion, migration and pollination, are influenced by more local circumstances (Morandin and Kremen 2013;Panagos et al. 2015;Shackelford et al. 2013;Wratten et al. 2012), the data for which are not available or suitable for this broad spatial analysis.
With respect to the EFAs, there are 19 that can be activated by Member States (MSs). Ten have been selected for inclusion in this study as they have the potential to affect the water-related ecosystem services selected. The EFAs are afforested areas, agroforestry, buffer strips, catch crops or green cover, ditches, fallow land, hedges or wooded strips, nitrogen fixing crops, ponds and short rotation coppice. The EFAs that have been excluded and their reasons for exclusion are: & Terraces: these only influence soil erosion in the indicator framework. & Isolated trees, field margins, stone walls and strips along forest edges: these do not influence the water-related ecosystem services in the indicator framework. Field margins could have an impact on water-related services, but in that instance they would be considered buffer strips, and thus are included in this study under that EFA. & Trees in line: the performance of this EFA in relation to water-related services is the same as hedgerows in the indicator framework, thus are included in this study under that EFA. & Trees in groups and field copses: the performance of this EFA in relation to water-related services is the same as afforested areas in the indicator framework, thus are included in this study under that EFA.

Data generation
The EFA calculator (AERU 2017; Tzilivakis et al. 2015b) is a standalone Microsoft Windowsbased software application that was originally designed to assess individual farms. A user enters data about the farm and its features that can be declared as EFAs, with the latter referring to the parcels of land (e.g. fallow land, catch crops, etc.) and landscape features (e.g. hedgerows, ditches, woodland, ponds, etc.). Each EFA is described in the software using quantitative dimensions (area, width, height, etc.) and a number of qualitative parameters (with classes within those parameters, e.g. soil texture is a parameter, with classes of coarse, medium, medium fine, fine and very fine). The underlying indicator framework (Tzilivakis et al. 2016) utilises these dimensions and parameter classes to assess the relative performance of each EFA with respect to its potential benefits and burdens on ecosystem services. Parameters and parameter classes have different weights and scores, respectively, which vary based on the relative significance of those factors for each EFA for each ecosystem service. Thus when each EFA is defined using these parameters, a score is derived for each ecosystem service. The output is a relative performance index (not quantified impacts or absolute values) on a scale of − 100 to + 100. Where data for some parameters are unknown, and thus unspecified, the software can calculate the worst, average and best case impacts for the feature, thus providing a potential range in impact.
Although the software is designed for use on individual farms, it has the potential to be used to support more strategic studies. For example, Angileri et al. (2017) used the tool to make an assessment of the potential impacts of EFA implementation at a regional level, by creating 121 hypothetical farms that were representative of a sample of NUTS3 regions across the EU (drawing upon data on the implementation of EFAs in those regions). A similar approach has been adopted in this study, except in this instance all NUTS3 regions have been assessed. However, running the EFA calculator software manually for all NUTS3 regions in the EU was not practical, therefore a bespoke batch processing routine was developed to automate the process. This included a parameterisation routine to automatically generate a farm for each region that has appropriate data for that region.
To create a farm for each NUTS3 region, the whole region was considered as a single farm. The size of the NUTS3 region and area of arable land in the region (sourced from EEA 2014) were used for the farm size and arable area respectively. Where the arable area for the region was zero, the region was excluded from the study. The data shown in Table 1 were used to derive region-specific parameter values for the farm. The EFA calculator software does account for more localised and/or management parameters, but these cannot be defined at a regional scale. The data for these parameters for each EFA were not set, i.e. were unspecified. Consequently, as described above, the known parameter values for each region in combination with the best and worst unspecified parameters were used to calculate worst, average and best case scenario values. Finally, to facilitate an individual analysis of each of the ten EFAs, a version of the farm was created to assess each EFA, with the area being set to 5% of the arable area. An example farm for Mittelburgenland in Austria (AT111) is shown in Table 2.
The process above resulted in 1256 NUTS3 farms, which were duplicated for each of the 10 EFAs, resulting in 12,560 files. These were then run through the EFA calculator twice, to generate a worst case and best case value for each impact, with the average case value calculated from these two values. Thus there were 37,680 sets of impact performance values output from the EFA calculator.

Data analysis
The data generated from the approach described in Section 2.2 needed to be combined with water-related ecosystem service vulnerability outputs from Tzilivakis et al. (2015a). In summary, these were:  The ecosystem service classification used by Tzilivakis et al. (2015a) is different to that used in the EFA calculator and indicator framework (Tzilivakis et al. 2016). The latter uses Version 4 of the Common International Classification of Ecosystem Services (CICES) system (Haines-Young and Potschin 2013), whereas the former uses a bespoke system. Therefore the classification of Tzilivakis et al. (2015a) was 'mapped' to the CICES classification in order to harmonise the two approaches and facilitate analysis as shown in Table 3 (Notes: (i) CICES uses a hierarchical classification, which is shown in Table 3; (ii) the latest version of CICES (Version 5.1) was not available at the time the study was undertaken. However, the extensions and revisions in the latest version do not impact upon the results presented in this study).
Deriving an assessment of the potential performance of EFAs in relation to the climate change vulnerabilities (Tzilivakis et al. 2015a) was undertaken in two stages. Firstly, the outputs from the EFA calculator were adapted using a weighting factor to generate a vulnerability weighted performance score for each EFA, for each ecosystem Where: Score VW Vulnerability weighted performance score Score Unweighted performance score for an EFA for an ecosystem service VC W Normalised vulnerability class weighting factor (see Eq. 2) The vulnerability classes were normalised on to a 0 to 100 scale using Eq. 2. The vulnerability classes needed a simple normalisation factor to convert them to a 0 to 100 scale. Where: VC W Normalised vulnerability class weighting factor VC Vulnerability class Nf Normalisation factor: the vulnerability classes derived by Tzilivakis et al. (2015a) have variable scales, e.g. 1-10 or 1 to 70, so required converting to a scale of 1 to 100 by applying a normalisation factor, e.g. flood regulation is 0 to 10, so a normalisation factor of 10 is applied to convert the class Those EFAs that have a high vulnerability weighted performance score are likely to be the most beneficial with respect to enhancing those ecosystem services in regions where they are most vulnerable to climate change. Water a Although a CICES class does exist for filtration (e.g. filtration/sequestration/storage/accumulation by ecosystems), the assessment of the performance of EFAs in the indicator framework (Tzilivakis et al. 2016) is more focused on the outcome, i.e. water quality in this instance. Hence filtration has been associated with the CICES chemical condition of freshwaters class The second stage accounts for the potential extent an EFA could be implemented within a region. This was done by using the percent arable area in a region to provide an area and vulnerability weighted performance score (Score VAW ) using Eq. 3. Where: Score VAW Vulnerability and area weighted performance score Score VW Vulnerability weighted performance score AA Percentage of arable area of the region (expressed as a fraction between 0 and 1) The above process resulted in 105,504 items of data (1256 NUTS3 regions × 2 impact values [positive and negative] × 3 scenarios [worst, average and best] × 14 EFA-ecosystem service combinations). It is not feasible, or particularly useful, to present this raw data in its entirety herein. Therefore to aid interpretation, the weighted performance scores were imported into a GIS compatible database and maps of NUTS3 regions were created using version 2.18 of QGIS (QGIS Development Team 2017). The coordinate reference system (CRS) used for the maps is ETRS89-LAEA Europe, also known in the EPSG Geodetic Parameter Dataset under the identifier: EPSG:3035. A worst, average and best case map has been created for each EFA-ecosystem service combination using the vulnerability and area weighted performance score (Score VAW ). The shading on the maps is red for burdens and green for benefits, with It is important to note that the numbers shown in Table 4 are the relative performance for the specific EFA only (i.e. not absolute values for the ecosystem services) and thus should not be used to compare one EFA to another. For example, a best case score of 16 for dilution for buffer strips is not equivalent to the score of 16 for dilution for ditches. It simply means they both have a moderate potential to contribute to dilution in their own specific way in regions where they achieve this score darker shades representing greater burdens or benefits. The gradient of the shading is based on the worst and best case values for each EFA for each ecosystem service (as shown in Table 4). Table 4 provides an overview of the worst and best unweighted and weighted performance scores for each EFA. The regional variability in the performance of the different EFAs for each ecosystem service is illustrated in the maps shown in Figs. 1, 2 , 3, 4, 5, 6, 7, 8, 9, 10, 11, 12, 13 and 14 (worst, average and best case scenarios from left to right) and main observations for each EFA have been drawn out in the discussion.

Interpretation and implications for EFA activation and implementation
This section explores the results of the spatial analysis with respect to countries and regions across Europe that have or have not activated each EFA. Table 5 provides an overview of which EFAs each MS has activated (note there are 32 as the UK and Belgium are split into 4 and 2 regions respectively) and Table 6 provides some example results for individual NUTS3 regions that are mentioned below.
Afforested areas The unweighted scores for afforested areas (Table 4) indicate that there are regions where the combination of attributes means that potential benefits and burdens are maximised (as indicated by the − 100 and + 100 scores). For dilution, the vulnerability (Score VW ) and area and vulnerability (Score VAW ) weighted scores are significantly lower, indicating that high vulnerability is not coinciding with the attributes for maximum impact and/or a high proportion of arable land in the region. This lack of coincidence is less so for flood regulation and water provision which have higher Score VW and Score VAW values. Thus it can be concluded that the implementation (or avoidance) of afforested areas has the greatest potential benefits with respect to flood regulation and burdens with respect to water provision, and lesser potential burdens with respect to dilution. The areas with the greatest potential benefits for flood regulation are those where the vulnerability to flooding is high, annual rainfall is high and there is a high proportion of arable land (thus high potential to implement this land use as an EFA). This includes central Denmark, eastern England, northwest France, central-northern Italy, central Greece, north-east Germany, southern Poland and Lithuania (see Fig. 1). There are some minor differences between the worst to best case scenarios. The areas with the greatest potential burdens for water provision are those where the region is vulnerable (i.e. currently water stressed and predicted to become warmer and drier) and paradoxically where rainfall is high (as there is greater scope for a reduction in water provision). This includes eastern-England, Denmark, northern France, central Spain, central Germany, Poland, eastern Italy, Hungary and southeast Romania (see Fig. 2). There are some major differences between the worst and best case scenarios, with the best case scenario eliminating any significant burdens, whilst the worst case scenario significantly extends the number of regions where burdens could occur. There are other more localised and management factors, which have not been specified in this spatial analysis, which affect the benefits and burdens (these unspecified factors contribute the difference between the worst and best case scenarios). These are that older woodlands (20+ years) tend to have a greater effect on flood regulation and water provision (Farley et al. 2005), with coniferous woodland having a slightly greater effect than broadleaved woodland (Sahin and Hall 1996).
The areas with the greatest potential burdens for dilution are those where vulnerability to dilution is high (i.e. where the current chemical condition of water is low, and the region is predicted to become drier resulting in less volume of water) and where the risk of acid and nutrient deposition is high and the buffering capacity of the soil is low. This includes include northern France and Belgium, eastern Spain, south and eastern Netherlands, western Germany, north and eastern Italy, Hungary and eastern Greece (see Fig. 3). There are some minor differences between the worst to best case scenarios. Other more geographically localised and/ or management factors that influence the burdens and were unspecified are woodland type (with coniferous and eucalypts having a greater burden than broadleaved woodland), and whether the woodland is commercially harvested or not, with commercially harvested woodlands having a slightly lower burden (Allen and Chapman 2001;Bastrup-Birk and Gundersen 2004).
There are eight MSs that have not activated the 'afforested areas' or the 'trees in groups and field copses' EFAs. Two of these have been identified as having significant potential for benefits for flood regulation (based on the combination of the performance of the EFA, the vulnerability and the area of arable land). These are (with example regions) Denmark (e.g. Sydjylland-DK032) and UK-England (e.g. Lincolnshire-UKF30). A further nine MSs have activated 'trees in groups and field copses' only, and two of these have been identified as having significant potential for benefits for flood regulation should there be more uptake of afforested areas. These are Greece (e.g. Larisa-EL612) and Lithuania (e.g. Siauliu apskritis-LT006).
It could be argued that these MSs should consider activating the 'afforested areas' EFA. However, there are also burdens from afforested areas on water provision and dilution. In many respects, this is a trade-off as the consequence of forests retaining water (to minimise flooding) is that this can reduce water provision and dilution downstream in the catchment. However, this trade-off depends on the circumstances of each region. With regard to water . Denmark and England, which could gain benefits for flood regulation by activating this EFA, also have areas that would experience significant burdens on water provision. Thus if activated, the potential trade-offs would need to be considered on a region by region basis. Potential dilution issues have been identified for Belgium, France, Germany, Italy, Spain which have activated 'afforested areas' and Greece and the Netherlands which have activated 'trees in groups and field copses' (e.g. Arr. Ieper-BE253, Somme-FR223, Emsland-DE949, Cremona-ITC4A, Teruel-ES242, Larisa-EL612 and Oost-Groningen-NL111). So again it may be advisable for these MSs to avoid implementing 'afforested areas' in regions most vulnerable to dilution issues, and Greece may also need to consider the trade-off between flood regulation benefits and dilution burdens on a region by region basis.
Agroforestry The unweighted scores for agroforestry (Table 4) indicate that there are no regions where the combination of attributes results in the potential benefits and burdens being maximised. The burdens are all very low and although there is some regional variation in the resulting burden (see Fig. 4), it is not significant enough to recommend the avoidance of implementing agroforestry to reduce burdens on dilution. where the combination of attributes means that the potential benefits for both dilution and filtration are high (as indicated by the + 78 score) and some regions where the combination of attributes results in low to moderate burden (− 15). The Score VW and Score VAW values are significantly lower for the burdens indicating that high vulnerability is not coinciding with the attributes for burdens and/or high proportion of arable land in the region. The benefits are also lower when weighted for vulnerability and area, but remain low to moderate (41 and 16 for dilution and 51 and 25 for filtration). Overall, this indicates there is scope for benefits from buffer strips and only a few locations where the burdens are likely to be minimal or negligible.
The areas with the greatest potential benefits for dilution and filtration from buffer strips include those where vulnerability to dilution and filtration are high, there is low annual rainfall, coarse soils and a high soil hydraulic conductivity for loss of phosphate and pesticides, moderate soil hydraulic conductivity for loss of nitrogen and there is a high proportion of arable land. For dilution (see Fig. 5), this includes northern France, and Belgium, eastern Spain, south and eastern Netherlands, western Germany, north-east and southern Italy, Hungary and eastern Greece. There are some minor differences between the worst and best case scenarios, but notably the worst case scenario results in some minor burdens in northwest Spain, northern Italy and central Germany. For filtration (see Fig. 6), there are very clear benefits in northern France, followed by southern England, northeast Italy and Hungary, with minor benefits across most other regions. In the main, differences between the worst and best case scenarios are minor, although the worst case scenario does result in some minor burdens France. Other more geographically localised and/or management factors that influence the benefits/burdens and were unspecified include the width of the buffer strip, vegetation height and density; slope; risk of overland flow becoming concentrated; removal of accumulated pollutants; erosion risk; presence of sub-surface drains; and the depth of impermeable layer beneath buffer strip (Bhattarai et al. 2009;Kay et al. 2009;Krutz et al. 2005;Reichenberger et al. 2007).
There are 15 MS that have not activated the 'buffer strips' EFA. Two of these have been identified as having significant potential for benefits for dilution, i.e. Czech Republic (e.g. Stredocesky kraj-CZ020) and Spain (e.g. Tarragona-ES514). Spain (e.g. Cádiz-ES612) and the Netherlands (e.g. West-Noord-Brabant-NL411) could also achieve minor benefits for filtration.
Catch crops or green cover The unweighted scores for catch crops or green cover (Table 4) indicate that there are regions where the combination of attributes results in moderate potential benefits for dilution (+ 36) and there are some regions where the worst case would result in a slight burden (− 6). The Score VW and Score VAW values are slightly lower for the best case scenario and significantly lower for the worst case scenario indicating that high vulnerability and/or a high proportion of arable land in the region, are only partially coinciding with the attributes for benefits and not coinciding for burdens. The areas with the greatest potential benefits for dilution from catch crops are those where the vulnerability to dilution is high and those which have coarse soils, high annual rainfall (i.e. those where leaching risk is high) and there is a high proportion of arable land. This includes Italy, northeast France, northern Belgium, western Germany, eastern and southwest Spain, Hungary and Greece (see Fig. 7). There are some minor differences between the worst and best case scenarios, with the worst case scenario resulting in minor burdens in northern France, northeast Spain, patches of central and eastern Germany, patches in Italy, Greece and Hungary. Other more geographically localised and/or management factors that influence the benefits/ burdens and were unspecified include slope, with flatter areas reducing the risk of losses via run-off and the catch crop species, with the greatest benefits provided by, for example, Brassica napus (rapeseed) and Hordeum vulgare (barley) and least by Zea spp. (maize) and Vicia sativa (common vetch) (depending on the other factors present) (Dabney et al. 2001;Novara et al. 2011;Ruiz-Colmenero et al. 2011;Shepherd 1999).
There are ten MSs that have not activated the 'catch crops or green cover' EFA. Three of these have been identified as having significant potential for benefits for dilution. These are Italy (e.g. Campobasso-ITF22), Spain (e.g. Cádiz-ES612) and Greece (e.g. Karditsa, Trikala-EL611).
Ditches The unweighted scores for ditches (Table 4) indicate that there are regions where the combination of attributes results in high potential benefit (+ 75) or moderate burden (− 20) for dilution, and the benefit is maximised (+ 100) for flood regulation. For dilution, the Score VW and Score VAW values are significantly lower indicating that high vulnerability and/or high proportion of arable land in the region are not coinciding with the attributes for high benefits or burdens, but they are still moderate and low for the best and worst case scenarios. For flood regulation, there is a greater coincidence with a maximum Score VW value (+ 100) and a slightly lower Score VAW value (+ 59). There is consequently scope for moderate to high benefits in relation to flood regulation, moderate benefits for dilution and low burdens for dilution.
The areas where ditches have a high benefit for flood regulation are simply those where the vulnerability to flooding is high and there is a high proportion of arable land. This includes central Denmark, eastern England, northwest France, central-northern Italy, central Greece, northeast Germany, southern Poland and Lithuania (see Fig. 8). There are some minor differences between the worst and best case scenarios, with the worst case scenario resulting in no benefits for flood regulation. Areas where ditches have benefits and burdens for dilution relate to the dilution vulnerability in the region and the proportion of arable land. The greatest benefits are in northern France and Belgium, eastern and southwest Spain, south and eastern Netherlands, western Germany, northeast and southern Italy, Hungary, southern Bulgaria and eastern Greece (see Fig. 9). There are some minor differences between the worst and best case scenarios, with the worst case scenario resulting in burdens in northern France, southeast England, eastern and southwest Spain, Germany, Czech Republic, Hungary, southern Romania, Bulgaria and Greece. The worst to best case scenarios are influenced by more geographically localised and/or management factors which have not been specified in this spatial analysis. These factors include disposal of cut weeds (whether they are removed or not), presence of low-grade weirs/small dams in ditch (with sediments removed periodically), the general in-ditch flow rate, the presence of in-ditch vegetation, dredging of ditch sediments, disposal of dredged sediments, time of dredging, whether high sulphate soil additions are used, intermittent periods of ditch drying and whether livestock have access to the ditch bank (Kröger et al. 2014;Needelman et al. 2007;Shore et al. 2015;Smith 2009).
There are 14 MSs that have not activated the 'ditches' EFA. Two of these have been identified as having significant potential for benefits for dilution. These are Spain (e.g. Cádiz-ES612) and Bulgaria (e.g. Yambol-BG343). Consequently, activation of this EFA in these regions may be beneficial. In the case of Bulgaria, the 'ditches' EFA was available in 2015-2016, but has been deactivated in 2017. The reasons for this are unknown, but it should perhaps be reconsidered for activation in the future. A number of MSs also have regions where low burdens in relation to dilution might result from ditches, such as Kilkis (EL523) in Greece.       However, it should be noted that the worst case values, as explained above, would only be realised under specific local and/or management factors. Two MSs that have not activated the 'ditches' EFA have been identified as having significant potential for benefits for flood regulation. These are Denmark (e.g. Sydjylland-DK032) and UK-England (e.g. Lincolnshire-UKF30).
Fallow land The unweighted scores for fallow land (Table 4) indicate that there are regions where the combination of attributes results in a moderate potential burden (− 36) for dilution. The Score VW and Score VAW values are lower indicating that high vulnerability and/or a high proportion of arable land in the region are not coinciding with the attributes for high burdens.
The areas with the greatest potential burdens for dilution from fallow land are those where the vulnerability to dilution is high, which have coarse soils, high annual rainfall (i.e. those where leaching or soil erosion risk is high) and where there is a high proportion of arable land. This includes northern France, eastern and southern Italy, Greece, Hungary, eastern and southwest Spain, central Germany and southern Bulgaria (see Fig. 10). There is only a small difference between the worst and best case scenario, with the best case having no burdens. Other more geographically localised and/or management factors which will affect the benefits/ burdens and were unspecified are ground cover and slope, with the worst case scenario being coarse soils, high rainfall, bare soil and steep slopes.
Only the Netherlands and Romania have not activated the 'fallow land' EFA. Under a worst case scenario, there is some potential for low burdens in both Romania (e.g. Teleorman-RO317) and the Netherlands (e.g. Zeeuwsch-Vlaanderen-NL341), but these are low values and thus are not sufficient to recommend avoiding fallow land (and with no benefits for dilution, there is no incentive activate this EFA) in these MSs.
For those MSs that have activated fallow land, northern France, eastern Italy and Greece and Hungary have regions where the worst case scenario could result in slightly higher burdens. For example, regions such as Somme (FR223), Ascoli Piceno (ITE34), Karditsa, Trikala (EL611) and Bekes (HU332) should perhaps avoid implementing fallow land with bare soil on steep slopes.
Hedges or wooded strips The unweighted scores for hedges or wooded strips (Table 4) indicate that there are regions where the combination of attributes results in a maximum potential benefit (+ 100) for dilution. The Score VW and Score VAW values are lower, but this relates to the vulnerability score and the proportion of arable land in the region. This includes northern France and Belgium, eastern and southwest Spain, south and eastern Netherlands, western Germany, northeast and southern Italy, Hungary and eastern Greece (see Fig. 11). There are some minor differences between the worst and best case scenarios, with the worst case scenario providing no benefits. The unspecified attributes that affect the performance of hedges with regard to dilution (other than vulnerability) are more localised and management factors, including the hedge height and porosity, whether pesticides are applied upwind and whether water bodies are downwind of the hedge (Hagen and Skidmore 1971;Rider 1952;Schwartz et al. 1995;Ucar and Hall 2001). These factors account for the range in performance from worst (0) to best case (21).
There are 13 MSs that have not activated the 'hedges or wooded strips' or 'trees in a line' EFAs. Two of these have been identified as having significant potential for benefits in relation to dilution. These are Spain (e.g. Cádiz-ES612) and Greece (e.g. Kilkis-EL523). In these countries, it is anticipated that trees in a line (i.e. shelterbelts) would be the EFA to be activated as hedgerows are a less traditional feature in these countries.
Nitrogen fixing crops The unweighted scores for nitrogen fixing crops (Table 4) indicate that there are regions where the combination of attributes results in a moderate potential burden for dilution (− 41). The Score VW and Score VAW values are lower indicating a high vulnerability and/or high proportion of arable land are not coinciding with the attributes for high burdens.
The areas with the greatest potential burdens for dilution from nitrogen fixing crops are those where the vulnerability to dilution is high, those which have coarse soils and high annual rainfall (i.e. those where leaching risk is high) and where there is a high proportion of arable land. This includes northern France, eastern and southern Italy, Greece, Hungary, eastern and southwest Spain, western Germany and southern Bulgaria (see Fig. 12). There is only a small difference between the worst and best case scenario, with the best case having no burdens. Other more geographically localised and/or management factors which will affect the benefit/burden and were unspecified are the crop species (which affects ground cover, and thus run-off and leaching losses) and slope, with the worst case scenario being coarse soils, high rainfall, steep slopes and species such as Galega spp. (Goat's rue), Pisum spp. (Pea), Vicia faba (Faba bean), Arachis spp. (Pinut) and Hedysarum coronarium (French honeysuckle) (Entrup and Stemann 1990;Jensen et al. 2010;Justus and Köpke 1995).
All MSs except for Denmark have activated the 'nitrogen fixing crops' EFA. There seems to be little scope for burdens in Denmark, so this EFA could be implemented for other benefits without incurring a burden in relation to dilution.
Ponds The unweighted scores for ponds (Table 4) indicate that there are regions where the combination of attributes results in a high potential benefit for dilution (+ 97). The Score VW and Score VAW values are significantly lower, but are still moderate (51 and 20). Overall, this indicates that there is scope for dilution benefits from ponds.
The areas with the greatest potential for benefits are those where the vulnerability to dilution is high, those which have a high annual temperature and there is a high proportion of arable land. This includes northern France, eastern and southern Italy, Greece, Hungary, eastern and southwest Spain, western Germany and southern Bulgaria (see Fig. 13). There is only a small difference between the worst and best case scenario, with the worst case having no benefits. Other more localised and management factors which will affect the benefit/burden and were unspecified are the pond size and average retention time, whether it is part of series of ponds and whether sediments are removed by dredging (Braskerud 2002a, b;Céréghino et al. 2014;IGER 2002;Ockenden et al. 2014).
Seventeen MSs have not activated the 'ponds' EFA. Three of these have been identified as having significant potential for benefits on dilution. These are Greece (e.g. Kilkis-EL523), Spain (e.g. Zaragosa-ES243) and Bulgaria (e.g. Yambol-BG343). Consequently, activation of this EFA in these regions may be beneficial. In the case of Bulgaria, the ponds EFA was available in 2015-2016, but has been deactivated in 2017. The reasons for this are unknown, but it should perhaps be considered for reactivation in the future.
Short rotation coppice The unweighted scores for short rotation coppice (Table 4) indicate that there are no regions where the combination of attributes means that potential benefits or burdens are maximised, there are just very low burdens. Although there are some regional variations within this slight burden (see Fig. 14), it is not significant enough to recommend the avoidance of implementing short rotation coppice to reduce dilution burdens.

Limitations and wider perspectives
This study has brought together the outputs from two continental-scale projects, both of which synthesised a substantial amount of scientific data and information. In some respects, it has been an exercise in the conversion of scientific knowledge into a format that can aid pragmatic decision making. This conversion process inherently involves aggregation and simplification and the application of novel processes and techniques. Consequently, it is important to acknowledge some of the weaknesses in the approach and any limitations on the findings of this study.
Firstly, it is important to acknowledge that the assessments have been made based on a knowledge base of existing evidence of the potential impact of EFAs, and this is not complete for all ecosystem services across all the EFAs. Consequently, there may be benefits and burdens for some ecosystem services from some of the EFAs explored in this study, which have not been highlighted in this analysis. For example, afforested areas are the only EFA that has been examined with respect to impacts on water provision. Other EFAs, such as agroforestry, ditches, hedges, ponds and short rotation coppice, may also have an impact. However, the knowledge base (Tzilivakis et al. 2015b) that underpins the indicator framework (Tzilivakis et al. 2016) is based on the weight of evidence that was available at the time, and there was a lack of scientific evidence specifically exploring the impact of these EFAs in relation to water provision. Similarly, only afforested areas and ditches have been examined with respect to impacts on flood regulation. Many other EFAs could also potentially affect hydrological processes and thus flood regulation, but again evidence associating (and quantifying) the effect of specific EFAs was lacking. This is not a new phenomenon, as all environmental assessments are made based on the most established and relevant scientific understanding available at the time. Scientific knowledge is evolving and growing all the time; consequently, efforts are ongoing to plug gaps in the knowledge base that underpins the EFA calculator, and as the science improves, the assessments made within the tool should reflect this.
It is important to acknowledge that the spatial analysis presented herein is a relatively broad-brush approach and that any benefits or burdens identified for a region do not mean this will definitely occur should those EFAs be implemented on any farm within the region. Specific benefits and burdens will depend on the details of their implementation on each farm within each region, e.g. buffer strips being located in the right places to be most effective in a catchment. The analysis presented herein does account for this to some extent by presenting the worst and best case scenarios (which account for unspecified parameters), but it is likely there will be greater variability.
In relation to the last point, it is also important to acknowledge that no account is taken of the performance of an EFA in a region in relation to a baseline. The analysis is simply highlighting the potential benefits and burdens should the EFA be implemented on 5% of the arable land within the region. The EFA policy only requires that an area of the farm that is equivalent to 5% of arable land area is declared as EFA. This may not necessarily require the creation of new EFAs, as EFAs covering 5% may already exist. The baseline situation could be accounted for within the spatial analysis by adjusting the area weighting using data on existing EFA declaration or using data such as the distribution of semi-natural vegetation in agricultural land (as done by Angileri et al. 2017). However, in this instance, the study is examining potential future vulnerabilities and the need to increase capacity within a region to cope with climate change. Therefore, the results presented herein should be interpreted as a need to increase certain EFAs in order gain the benefits (or avoiding certain EFAs to decrease burdens).
It is also important to reiterate that the indicator framework used (Tzilivakis et al. 2016), and thus the analysis presented, is one that identifies the relative performance of an EFA and does not quantify actual benefits or burdens for ecosystem services. Quantification of ecosystem services requires more sophisticated techniques, many of which do not exist for such broad-scale analyses (Baveye 2017;Maes et al. 2016). Efforts are being made to develop such techniques, such as those that have emerged from the Quantification of Ecological Services for Sustainable Agriculture project (QuESSA 2017). Some of these have been incorporated into the latest version of the EFA calculator, but these are only available for a limited number of ecosystem services, including pollination, pest control, soil erosion, carbon and aesthetics. As such techniques evolve and develop, a similar analysis to the one presented herein could be undertaken using these techniques, and could liberate additional information that could aid decision making and the selection and implementation of EFAs that maximise benefits and minimise burdens for ecosystem services under current and future climatic scenarios.
This study has explored the potential benefits and burdens of EFAs on water-related ecosystem services vulnerable to climate change. It is important to remember that the EFAs examined in this study (and those not examined) also have other benefits and burdens which will influence decisions with regard to their promotion (via policy) and uptake on the ground. There can be numerous effects and impacts to consider, for example climate regulation (greenhouse gas emissions, including above and below ground carbon), soil erosion, pollination, pest control, aesthetic and other cultural services and biodiversity. Some of these could be explored using the spatial analysis presented herein, but many will depend on more localised variables and management factors for which georeferenced spatial data do not exist. Should this data for these factors become available, then these could be analysed in the same way, extending the assessment to include more ecosystem services and EFAs, and thus providing a more holistic perspective.
It is important that other benefits and burdens are taken into account in the decision making processes associated with their promotion, uptake and implementation. This will involve identifying where there are synergies and trade-offs to be taken into account. The spatial analysis presented in this study can support these decision making processes by identifying regions where the greatest benefits and burdens might occur in the event of climate change projections being realised. For example, afforested areas have the potential to provide benefits for flood regulation and burdens for water provision and dilution. Under the right circumstances, they can also provide benefits for numerous wildlife species, climate regulation (via carbon sequestration), pollination and aesthetic services. The synergies and trade-offs between these benefits and burdens will need to be considered within each region when considering the implementation of EFAs. As such, the spatial analysis presented herein can contribute towards understanding such synergies and trade-offs in the context of future vulnerabilities and threats from climate change.
This study has explored the potential impact on ecosystem services from a number of land uses and landscape features in the context of Europe and its land use policies in the light of projected changes in climate in the future. Other continents and countries around the world face similar challenges (Chang and Bonnette 2016;Fu et al. 2017;Malinga et al. 2015;Overbeck et al. 2015;Rodríguez-Echeverry et al. 2018;Tolessa et al. 2017), so there is a need for tools and techniques to aid policy assessment and development. For example, Tolessa et al. (2017) utilised GIS techniques to estimate changes in ecosystem services over 40-year period as a consequence of land use change in the central highlands of Ethiopia. This study highlighted the impact of Ethiopian land use policies during this period and thus can be used to adapt policies towards sustaining important ecosystem services. Similarly, Rodríguez-Echeverry et al. (2018) adopted a spatial approach to assess the impact of land use change ecosystem services from Chilean temperate forests and identified that losses in habitat and diversity are having detrimental effects on soil erosion and water supply. Fu et al. (2017) also used a spatial approach to assess the effects of land use and climate change on ecosystem services in central Asia's arid regions and propose a number of policy responses to sustain ecosystem services. All these studies attempt to take into account land use, ecosystem service provision and vulnerability to climate change. An important element amongst them all is the utilisation and tailoring of appropriate measures and indicators in the regions being studied. The study presented herein demonstrates how an indicator framework can be developed based on the latest knowledge of the effects and impacts of land use and then applied in the context of climate change vulnerability using spatial techniques. This 'generic' concept could be applied elsewhere in the world and thus help spatially target mitigation and adaptation policy interventions based on current knowledge and understanding in any given region.

Conclusions
There is little doubt that climate change and its consequent effects and impacts pose a great challenge to society, thus there is a need for robust mitigation and adaptation strategies and policies. Understanding the threats and vulnerabilities is a key aspect to tackle this challenge.
Another key aspect is to determine the actions that will minimise any negative effects and impacts. This applies to all industry sectors, including rural land management, and applies to both policy makers and managers on the ground. It is important that relevant stakeholders have access to reliable information, data and analysis that will aid decision making on what are often complex topics. This often involves processing a substantial amount of complex data and information and presenting and interpreting it in a form to support decision making processes.
This study has used the continent of Europe as example to explore the challenges involved in assessing the benefits and burdens of land use policies on water-related ecosystem services that are vulnerable to climate change. Many of these are common to other regions of the world, for example water provision/supply in California, USA (Byrd et al. 2015), Chile (Rodríguez-Echeverry et al. 2018) and Ethiopia (Tolessa et al. 2017); water regulation and flooding in China (Ouyang et al. 2016) and the USA (Blumstein and Thompson 2015); and water quality in China (Gao et al. 2017) and Japan (Fan and Shibata 2015). Consequently, the study presented in this paper has global relevance. Many of the land uses and landscape features explored in this study exist in other regions of the world. The effects and impacts will vary with location, as they do in Europe, but under similar circumstances, similar benefits and burdens may arise. Where circumstances are different, the approach presented in this paper of combining pertinent indicators, spatial data and vulnerability assessments could be applied to other regions and continents to aid the development of mitigation and adaptation strategies and policies for land use and ecosystem services.
This study combined the outputs from two continental-scale projects to provide a means to identify European regions where EFAs may help increase the capacity of water-related ecosystem services in areas where they are vulnerable due to climate change. Six EFAs have been identified which have not been activated in some MSs, but which have the potential to provide benefits. These include afforested areas for flood regulation in Denmark, England, Greece and Lithuania; buffer strips for dilution and filtration in the Czech Republic, Netherlands and Spain; catch crops or green cover for dilution in Greece, Italy and Spain; ditches for dilution in Bulgaria and Spain and for flood regulation in Denmark and England; trees in a line (hedges) for dilution in Greece and Spain; and ponds for dilution in Bulgaria, Greece and Spain. It is recommended that these MSs consider activating these EFAs in the future. Eleven Member States have also been identified which have regions where some EFAs should perhaps be avoided, due to potential burdens on vulnerable ecosystem services. These include afforested areas for water provision in some regions in France, Germany, Hungary, Italy, Poland, Romania and Spain, and for dilution in some regions in Belgium, France, Germany, Italy, Spain, Greece and the Netherlands; fallow land for dilution in some regions in the Netherlands, Romania, France, Italy, Greece and Hungary; and nitrogen fixing crops for dilution in some regions in Bulgaria, France, Germany, Greece, Hungary, Italy and Spain.
Current European policy does not require that new EFAs be created to meet the 5% arable area threshold for farms, as existing land use and landscape features can be declared as EFAs. This is still a positive policy as it aims to maintain these areas for the future. However, given the challenges that lie ahead with respect to climate change, there is a growing need to increase, rather than just maintain, the capacity of landscapes to perform the ecosystem services that society relies on, such as water provision, flood regulation and the water purifying services of filtration and dilution. As such, EFAs and/or other land management policies need to encourage this increase in capacity, especially in the most vulnerable regions.
It will also be important to ensure that there are demonstrable benefits from the implementation of EFAs or other interventions. The impact of land use policies on ecosystem services should be monitored to ensure expected outcomes are realised, and when they are not realised evidence on the reasons for this should be gathered. This will generate new scientific data, evidence and understanding that can be used to improve the knowledge base, improve the tools available to aid future decision making and consequently make progress towards more sustainable and resilient land use that delivers the ecosystem services society requires.